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MDBA Publication No: 28/12
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Title:
Assessment of environmental water requirements for the proposed Basin Plan:
Macquarie Marshes
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Macquarie-Castlereagh Region
Assessment of Macquarie Marshes environmental water
requirements
1. Introduction
The Water Act 2007 (Cwlth) established the Murray‐Darling Basin Authority (MDBA) and tasked it
with the preparation of a Basin Plan to provide for the integrated management of the Basin’s water
resources. One of the key requirements of the Basin Plan is to establish environmentally sustainable
limits on the quantities of surface water that may be taken for consumptive use, termed Sustainable
Diversion Limits (SDLs). SDLs are the maximum long‐term annual average volumes of water that can
be taken from the Basin and they must represent an Environmentally Sustainable Level of Take
(ESLT).
The method used to determine the ESLT is described in detail within ‘The proposed “environmentally
sustainable level of take” for surface water of the Murray-Darling Basin: Method and Outcomes,’
(MDBA 2011). A summary of the main steps undertaken to determine the ESLT is presented in
Figure 1. The assessment of environmental water requirements including specification of sitespecific flow indicators at a subset of hydrologic indicator sites (Step 3 of the overall ESLT method) is
the focus of this document.
The work described herein is the MDBA’s current understanding of the environmental water
requirements of the Macquarie Marshes. It is not expected that the environmental water
requirements assessments will remain static, rather it is intended that they will evolve over time in
response to new knowledge or implementation of environmental watering actions. Within this
context, feedback is sought on the material presented within this document whether that be as part
of the formal draft Basin Plan consultation phase or during the environmental watering
implementation phase within the framework of the Environmental Watering Plan.
1.1. Method to determine site-specific flow indicators
Assessment of environmental water requirements for different elements of the flow regime using
the hydrologic indicator site approach is one of the key lines of evidence that has informed the
proposed SDLs. Effort focussed on regions and parts of the flow regime with greatest sensitivity to
the scale of reduction in diversions necessary to achieve environmental objectives, an ESLT and a
healthy working Basin.
Within the overall framework of the ESLT method (Figure 1) the MDBA used an iterative process to
assess environmental water requirements and develop site-specific flow indicators.
The hydrologic indicator site approach uses detailed eco-hydrological assessment of environmental
water requirements for a subset of the key environmental assets and key ecosystem functions
across the Basin. Effort focused on high flow (freshes, bankfull flows and overbank flows)
requirements reflecting the prioritisation of effort on parts of the flow regime that are most
sensitive to the determination of the ESLT and SDLs. The Macquarie Marshes is one of the key
1
environmental assets where a detailed assessment of environmental water requirements was
undertaken.
Detailed environmental water requirement assessments lead to the specification of site-specific flow
indicators to achieve site-specific ecological targets. Flow indicators were expressed at a hydrologic
indicator site or sites. Environmental water requirements specified at hydrologic indicator sites are
intended to represent the broader environmental flow needs of river valleys or reaches and thus the
needs of a broader suite of ecological assets and functions.
Figure 1: Outline of method used to determine an Environmentally Sustainable Level of Take.
(Source: MDBA 2011).
This report provides a description of the detailed eco-hydrological assessment of environmental
water requirements for the Macquarie Marshes including information supporting the development
2
of site-specific flow indicators for the site (with reference to flows gauged on the Macquarie River at
Marebone Weir). More information on how the site-specific flow indicators for the Macquarie
Marshes were used within the Basin-wide modelling process to inform the ESLT (i.e. Step 5 and 6 in
Figure 1) can be found in the report ‘Hydrologic modelling to inform the proposed Basin Plan:
Methods and results’ (MDBA 2012).
A description of the detailed eco-hydrological assessments of environmental water requirements for
other indicator sites are described in other documents in the series ‘Assessment of environmental
water requirements for the proposed Basin Plan’.
1.2. Scope and purpose for setting site-specific flow indicators
The MDBA’s assessment of environmental water requirements and associated site-specific flow
indicators at hydrologic indicator sites has been used to inform the development of SDLs. This
enables the MDBA to estimate the amount of water that will be required by the environment over
the long-term to achieve a healthy working Basin through the use of hydrological models.
Accordingly, site-specific flow indicators are not intended to stipulate future use of environmental
water. MDBA expects that the body of work undertaken to establish these site-specific flow
indicators will provide valuable input to environmental watering but this watering will be a flexible
and adaptive process guided by the framework of the Environmental Watering Plan and natural ecohydrological cues. It will be up to the managers of environmental water, such as the Commonwealth
Environmental Water Holder, State Government agencies, and local communities to decide how best
to use the available environmental water during any one year to achieve environmental outcomes.
2. Site location and extent
The Macquarie Marshes hydrologic indicator site is an extensive wetland system on the lower
reaches of the Macquarie River in central New South Wales. The Marshes begin downstream of
Warren and extend about 120 km to near Carinda (NSW Department of Water Resources 1991), as
shown in Figure 2.
The Macquarie Marshes cover about 200,000 ha and include areas inundated by flows from the
Macquarie River and its streams and anabranches, specifically the Macquarie River, Marebone
Break, Bulgeraga Creek, Buckiinguy Creek, Monkeygar Creek, Old Macquarie River, Bora Channel, the
Ginghet, Mullins Swamp, Gum Cowal – Terrigal Creek to its confluence with Marthaguy Creek, Long
Plain Cowal and Dusty Swamp (NSW Department of Water Resources & NSW National Parks and
Wildlife Service 1986; NSW National Parks and Wildlife Service & Department of Land and Water
Conservation 1996; NSW Department of Environment, Climate Change and Water 2010a).
Most of the Marshes are privately owned, except for about 22,300 ha managed by the NSW Office of
Environment and Heritage, which includes the Macquarie Marshes Nature Reserve and the property
Pillicawarrina (NSW Department of Environment, Climate Change and Water 2010a; NSW
Department of Environment, Climate Change and Water 2010b). The Macquarie Marshes Ramsar
sites covers 18,726 ha and include the Macquarie Marshes Nature Reserve as well as the privately
owned Wilgara Wetland and Mole Marsh (Department of the Environment, Water, Heritage and the
Arts 2010). The Nature Reserve and Mole Marsh were listed as Ramsar sites in 1986 and the Wilgara
Wetland was listed in 2000 (NSW Department of Environment, Climate Change and Water 2010a;
3
Department of the Environment, Water, Heritage and the Arts 2010). Recently the property Ninia
was added to the Nature Reserve (Figure 2).
Figure 2 Location and extent of Macquarie Marshes hydrologic indicator asset
4
Generally the Marshes are subdivided into the Southern Marsh starting from near Marebone to
Mole Marsh, the Northern Marsh from Mole Marsh north along the Macquarie River and Bora Creek
system to near Carinda, and the East Marsh along the Gum Cowal Creek system (Figure 2) (NSW
Department of Environment, Climate Change and Water 2010c).
The Murray–Darling Basin Authority (MDBA) used the Directory of important wetlands in Australia
dataset (Department of the Environment, Water, Heritage and the Arts 2001) to map the lateral and
longitudinal extents of the Macquarie Marshes. The Ramsar Wetlands in Australia dataset was used
to define the western extent of the system. Spatial data used in this map is listed in Appendix A.
3. Ecological Values
The Marshes support a variety of flood-dependent vegetation types that include extensive water
couch (Paspalum distichum) and common reed (Phragmites australis) grasslands, river red gum
(Eucalyptus camaldulensis) forest and woodland, coolibah (E. coolabah) and black box
(E. largiflorens) woodland, and lignum (Muehlenbeckia florulenta) and river cooba (Acacia
stenophylla) shrublands (Paijmans 1981; Bowen and Simpson 2009). They are an important example
of associations of these vegetation types (NSW National Parks and Wildlife Service 1993;
Department of the Environment, Water, Heritage and the Arts 2010).
Species and communities that do not depend on flooding to complete their life cycle occur on the
edge of flooded areas and as pockets within the Marshes. These areas are flooded rarely or not at
all, and include weeping myall (A. pendula), belah (Casuarina cristata), and poplar box (E. populnea)
woodlands, chenopod shrublands, and grasslands (Paijmans 1981; Bowen and Simpson 2009).
Extensive areas of common reed and water couch and stands of cumbungi (Typha domingensis and
Typha orientalis) provide critical habitat for waterbirds and other wetland animals in the Marshes
(NSW Department of Environment, Climate Change and Water 2010c). Much of the 19,000 ha that
supported these communities in 1991 no longer contains flood-dependent vegetation. More than
half has been replaced by chenopod shrubland (Wilson 1992; Bowen and Simpson 2009).
River red gum forests and woodlands are also a distinctive feature of the Marshes. They are among
the most diverse of the wetland communities in the Marshes, and many have an understorey of
aquatic species (Bowen and Simpson 2009; NSW Department of Environment and Climate Change
2009a). River red gum provides critical habitat for waterbirds and other wetland animals, and is the
tree species most used for nesting by colonial nesting waterbirds in the Marshes (Oliver and Parker
2006; Blackwood et al. 2010).
Lignum and river cooba shrubland and coolibah and black box woodland are also important flooddependent species in the Marshes, providing critical habitat for many birds and animals (NSW
Department of Environment, Climate Change and Water 2010c). Lignum occurs in areas flooded at
frequencies of once in 2 to 10 years for durations of 3 to 12 months (Roberts and Marston 2011).
Found throughout the Marshes as an understorey plant, lignum provides critical breeding habitat for
waterbirds, especially ibis species.
5
Black box is found in the Marshes on less frequently flooded parts of the floodplain where it forms
black box and coolibah – black box woodlands. Coolibah – black box woodland is listed as an
endangered ecological community under the NSW Threatened Species Conservation Act 1995 (NSW
Department of Environment and Climate Change 2009a).
The Macquarie Marshes are one of the more important wetlands in Australia for breeding of colonial
nesting waterbirds (Kingsford and Auld 2005). Seventy-six waterbird species have been recorded in
the Marshes, 42 of which have been recorded breeding. Species include some listed as being
threatened both in New South Wales and nationally, as well as the only recorded pied heron (Ardea
picata) breeding in New South Wales (NSW Department of Environment, Climate Change and Water
2010c). Sixteen species have been recorded breeding, with the eastern great egret (A. modesta),
intermediate egret (A. intermedia), little egret (Egretta garzetta), rufous night heron (Nycticorax
caledonicus), glossy ibis (Plegadis falcinellus), Australian white ibis (Threskiornis molucca), strawnecked ibis (T. spinicollis), little pied cormorant (Phalacrocorax melanoleucos) and little black
cormorant (P. sulcirostris) occurring in the largest numbers (Kingsford and Johnson 1998; Kingsford
and Auld 2005). Most breeding sites are located in semi-permanent wetland vegetation and river red
gum forest and woodland, requiring frequent and prolonged flooding (Kingsford and Auld 2005;
NSW Department of Environment, Climate Change and Water 2010c).
The Macquarie Marshes have long been regarded as an important refuge for waterbirds during dry
times, as well as supporting some of Australia’s largest recorded waterbird breeding colonies
(Macquarie Marshes Investigation Committee 1951; Marchant and Higgins 1990; Kingsford and
Johnson 1998; Kingsford and Auld 2005).
The Macquarie Marshes support many important species that are listed in international agreements
and include vulnerable and endangered species. Appendix B provides a summary of the
conservationally significant species recorded at the site.
The ecological value of Macquarie Marshes is reflected in its rating against the criteria used by the
MDBA to identify key environmental assets within the Basin. The MDBA established five criteria
based on international agreements and broad alignment with the National Framework and Guidance
for Describing the Ecological Character of Australian Ramsar Wetlands (Department of the
Environment, Water, Heritage and the Arts 2008) and the draft criteria for identifying High
Conservation Value Aquatic Ecosystems (SKM 2007). Based on the ecological values identified at the
Macquarie Marshes, the site meets all of the five criteria for determining a key environmental asset
(Table 1).
6
Table 1 Assessment of the Macquarie Marshes against MDBA key environmental asset criteria
Criterion
Ecological values that support the criterion
1. The water-dependent
The Macquarie Marshes are formally recognised in, or are capable of supporting species
ecosystem is formally
listed in the Japan–Australia, China–Australia or Republic of Korea – Australia migratory
recognised in
bird agreements. The Macquarie Marshes Nature Reserve, Mole Marsh and the Wilgara
international agreements
Wetlands met the five criteria for Ramsar listing.
or, with environmental
watering, is capable of
supporting species listed
Species listed in international agreements that have been recorded at Macquarie Marshes
are in Appendix B.
in those agreements
2. The water-dependent
The Macquarie Marshes are one of the largest inland semi-permanent wetlands in south-
ecosystem is natural or
east Australia. The site is rare in terms of both its size and diversity of wetland types
near-natural, rare or
(Paijmans 1981; NSW National Parks and Wildlife Service1993; NSW Department of
unique
Environment, Climate
The
Change
water-dependent
and Water 2010c).
ecosystem is natural or near-natural, rare or unique
3. The water-dependent
The Macquarie Marshes are renowned for supporting large waterbird breeding events. The
ecosystem provides vital
Marshes are one of the few places in Australia that support large breeding colonies of
habitat
straw-necked ibis, asThe
wellwater-dependent
as some of the largest
ecosystem
breeding
provides
colonies
vital habitat
of intermediate egret,
rufous night heron and royal spoonbill (Platalea regia) in southern Australia. Many other
waterbirds, including cormorants, herons and ducks, also breed there. The Marshes are
one of the few sites in New South Wales where magpie geese (Anseranas semipalmata)
breed (Kingsford and Auld 2005; NSW Department of Environment and Climate Change
2006; Department of Environment, Climate Change and Water 2010b). These remaining
wetlands have become a regionally important refuge for wildlife, and an important drought
refuge.
4. Water-dependent
ecosystem that supports
Species and communities listed as threatened under both Commonwealth and state
legislation that have been recorded at the site are listed in Appendix B..
Commonwealth, state or
territory listed threatened
species or communities
5. The water-dependent
Water-dependent ecosystem that supports Commonwealth, state or territory listed threatene
The Macquarie Marshes support significant biodiversity (NSW National Parks and Wildlife
ecosystem supports, or
Service 1993; NSW Department of Environment, Climate Change and Water 2010c). They
with environmental
regularly support more than 20,000 waterbirds and over 500,000 waterbirds in large
watering is capable of
floods, including substantial numbers of cormorants, herons, ibises, spoonbills, swans,
supporting, significant
geese, ducks, raptors and migratory waders (Department of the Environment, Water,
biodiversity
Heritage and the ArtsThe
2010).
water-dependent ecosystem supports, or with environmental watering, is capable of sup
7
4. Hydrology
The Macquarie River rises on the western side of the Great Dividing Range, south-east of Bathurst,
and flows about 500 km north-west and north before joining the Barwon–Darling River in northern
New South Wales. The main tributaries enter the river upstream of Narromine and most are
upstream of Burrendong Dam, the river’s largest water storage. As the Macquarie flows onto the
Darling riverine plain downstream of Narromine, it develops distributary streams and forms
extensive floodplain wetlands (NSW Department of Water Resources 1991). These streams flow
north and north-west to join the Bogan and Barwon Rivers. The main Macquarie River channel
continues north from Narromine, forming the Macquarie Marshes about 50 km north of Warren.
The Marshes extend for about 120 km to Carinda before the river re-forms and flows to the Barwon
River between Walgett and Brewarrina (NSW Department of Water Resources 1991).
The upper Macquarie catchment has winter-dominant rainfall of between 600 mm and 1,000 mm
per year and evaporation of about 1,300 mm/y. The climate of the lower Macquarie is hot and semiarid, with summer-dominant rainfall averaging about 400 mm/y and evaporation of about
2,000 mm/y.
Most of the river flow comes from rainfall in the catchments upstream of Narromine. Annual flows
in the Macquarie River are extremely variable. Recorded flows at Dubbo range from 2% to 900% of
average flow since records were first kept in 1898 (NSW Department of Water Resources 1991).
Studies using measured and modelled flow data have found significant changes to the flow regime of
the river due to river regulation and extraction, including:





reduced moderate-to-high flows in the Macquarie River and end-of-system flows (CSIRO
2008);
an increase in the average period between large flows exceeding 200 GL volume between 1
June to 30 November at the Oxley gauge by 114% or from 2.2 years to 4.7 years on average
and a reduction in the average volume of these events, from 328 GL to 278 GL per event
(CSIRO 2008);
a reduction in the number of small flows greater than 1 GL/d likely to cause flooding passing
the Oxley gauge since construction of Burrendong Dam (Jenkins and Wolfenden 2006, in
NSW Department of Environment and Climate Change 2009a);
permanent low flows in previously intermittent streams (Grimes 2001); and
a significant reduction in the frequency of floods in the Marshes and the area inundated
(Thomas et al., in prep. (b); NSW Department of Environment and Climate Change 2009a).
5. Determining the site-specific flow indicators for the Macquarie
Marshes
5.1. Setting site-specific ecological targets
The objective setting framework used to determine the ESLT is outlined in the report ‘The proposed
“environmentally sustainable level of take” for surface water of the Murray-Darling Basin: Method
8
and Outcomes’ (MDBA 2011). In summary, the MDBA developed a set of Basin-wide environmental
objectives and ecological targets, which were then applied at a finer scale to develop site-specific
objectives for individual key environmental assets. Using these site-specific objectives, ecological
targets that relate specifically to the Macquarie Marshes were developed (Table 2). Information
underpinning site-specific ecological targets is shown in Table 2.
Site-specific ecological targets formed the basis of an assessment of environmental water
requirements and the subsequent determination of site-specific flow indicators for the Macquarie
Marshes, as described below.
Table 2 Site-specific ecological targets for Macquarie Marshes
Site-specific ecological targets
Justification of targets
 Provide a flow regime which supports
the habitat requirements of
waterbirds and is conducive to
successful breeding of colonial
nesting waterbirds
To breed successfully, colonial nesting waterbirds require, at a minimum,
flooding of sufficient volume and duration for colony sites and feeding areas
to be inundated for at least four to five months between August and March
(NSW Department of Environment, Climate Change and Water 2010c).
These flows are also critical for maintaining wetland vegetation and to
complete aquatic invertebrate life cycles (Jenkins and Wolfenden 2006).
 Provide a flow regime which ensures
the current extent of native
vegetation of the riparian, floodplain
and wetland communities is
sustained in a healthy, dynamic and
resilient condition
Wetland vegetation is the critical component that provides both diversity and
waterbird habitat.
 Provide a flow regime which supports
recruitment opportunities for a range
of native aquatic species (e.g. fish,
frogs, turtles and invertebrates)
 Provide a flow regime which supports
key ecosystem functions, particularly
those related to connectivity between
the river and the floodplain
It is highly likely that insufficient flow size, frequency, duration and timing will
cause a decline in the health of wetland vegetation, waterbird habitat,
aquatic ecology and waterbird breeding sites at the Macquarie Marshes
Nature Reserve Ramsar site. Threats associated with water availability and
water management are applicable to both this Ramsar site and the entire
Macquarie Marshes (NSW Department of Environment and Climate Change
2009b).
Bowen and Simpson (2009) outline changes in extent and condition of the
vegetation communities of the Macquarie Marshes in the period 1991–2008.
This information has been used as a basis for the vegetation targets.
Given the extent of changes to the hydrology and ecology of the Macquarie
Marshes, maintaining the extent of flood-dependent vegetation communities
at 1991 levels is considered to be unachievable through the Basin Plan.
5.2. Determining site-specific flow indicators
The following sections outline the various lines of evidence (e.g. ecological, hydrological and
geomorphological) and the method used to determine the environmental watering requirements of
the Macquarie Marshes to meet the site-specific ecological targets in Table 2.
5.2.1
Wetlands and vegetation
The ecological targets for the site are not aimed at restoring all flood-dependent vegetation
communities to their previous extent. Many areas of the Marshes no longer support wetland
vegetation. Erosion and channel formation mean it will not be possible to return flows to many areas
without substantial structural works. The nature and extent of these works is beyond the scope of
the Basin Plan.
9
For example, in 1991 about 39,000 ha of river red gum forest and woodland were mapped in the
Marshes (Wilson 1992). The condition of large areas of this forest and woodland has changed since
1991 because of changes in flow regime. Most areas now have an understorey dominated by
chenopod shrubs (Bowen and Simpson 2009; NSW Department of Environment and Climate Change
2009a). Many areas show a significant decline in canopy condition, with more than half the area
mapped in 1991 recently showing more than 40% dead canopy (Bowen and Simpson 2009).
Restoration of the extent of river red gum forest and woodland to the extent recorded in 1991 is
considered unachievable.
The main flood dependant vegetation types of the Macquarie Marshes are described in Bowen and
Simpson (2009), and summarised above in Section 3. These vegetation types require different
watering regimes. Roberts and Marston (2011) provides the most up-to-date information on
watering requirements of flood dependant vegetation species in the Murray–Darling Basin. Based on
this work, water requirements for the flood-dependent vegetation communities of the Macquarie
Marshes are shown in Table 3.
The NSW Department of Environment, Climate Change and Water (2010c) analysed historical
inundation patterns of the Macquarie Marshes, linking the inundation extent of historical flow
events to river flow data at Marebone Weir. This work provides an understanding of the flows
required to achieve different levels of inundation. Based on this analysis, the MDBA selected the
following flow events (volumes) to represent the typical range of environmental watering events
(from small to large) in the Macquarie Marshes; 100 GL, 250 GL, 400 GL, 700 GL and 1,300 GL. These
volumes are measured over 5 successive months June to April/May.
To gain an understanding of the frequency of these events, and an indication of the potential
associated outcomes, the MDBA assessed modelled without-development flow data for the period
1895 to 2009. This analysis showed that events of 1,300 GL volume are relatively rare, occurring in
only 3% of years under without-development conditions. Current understanding of the water
requirements of flood dependant species (e.g. Roberts and Marston 2011) indicates that events of
this frequency are unlikely to be critical to support flood-dependent vegetation. The extremities of
the floodplain, watered by large, infrequent events of this size, are likely to support flood tolerant
vegetation communities that are more dependent on local rainfall or groundwater for their survival.
Consequently, the MDBA used the 100GL, 250 GL, 400GL and 700 GL flood events as flow indicators
for the Macquarie Marshes.
A comparison of inundation extents with vegetation mapping undertaken by Bowen and Simpson
(2009) in 2008 enabled the proportions of vegetation communities inundated by the specified flow
volumes to be estimated. Table 4 has been adapted from NSW Department of Environment, Climate
Change and Water (2010c) and shows the area of key flood-dependent vegetation estimated to be
inundated by the selected flow volumes.
10
Table 3 Water requirements of vegetation communities in the Macquarie Marshes (adapted from Roberts and Marston 2011).
Species
Maintenance
Regeneration
Critical interval
Flood frequency
Flood duration
Timing of flooding
Black box
(Eucalyptus
largiflorens)
1 in 3- 7 years
3-6 months for vigorous canopy and
flowering. 2-3 months for moderate
to good canopy and flowering.
Tolerates shorter flooding, but
becomes less vigorous.
Probably not
important.
Advisable to follow
natural timing for a
site, where known
Germination on wet soils on flood
recession or in run on areas after rain.
Spring-Summer recession favours
seedling growth.
Re-flooding 3-7 years to maintain good
condition. Trees may survive 12-16 years
with no flooding but in poor condition,
forming dysfunctional woodlands, and with
diminished capacity for full recovery.
River red gum
(Eucalyptus
camaldulensis)
forests
1 in 1-3 years
5-7 months. Individual floods may
be longer or shorter without major
consequence; some variability is
encouraged.
Not critical. More
growth achieved in
spring and summer
More growth after spring-summer
floods. Warm, moist soil conditions best
for germination and seeding growth.
Flooding for 4-6 weeks duration is
adequate for re-generation.
Reflood after about 3 years if trees are to
retain vigour. Longer intervals may be
tolerated periodically, but if these become
routine tree condition is likely to deteriorate
in long term.
River red gum
woodlands
1 in 2-4 years
2-4 months. Individual floods may
be longer or shorter without major
consequence; some variability is
encouraged.
As for river red gum
forests
As for river red gum forests
Reflood after about 5-7 years if trees are
to retain vigour. Longer intervals may be
tolerated, but if these become routine tree
condition likely to deteriorate in long term.
Lignum
(Muehlenbeckia
florulenta)
1 in 1-3 years for
large shrubs
3-7 months for vigorous canopy
Not critical
Sequential or sustained flooding may
be needed to trigger flowering, set and
disperse seeds. Brief follow-up flooding
in 9-12 months increases seedling
establishment but not critical.
Reflood after 5-7 years to maintain vigour.
Rootstock may survive unflooded for up to
10 years, but branches totally dead. Must
be followed by optimal flooding conditions
to re-establish vigour.
River oak
(Casuarina
cunninghamiana)
In-channel freshes and overbank flows provide the flow variability that is
probably important in maintaining groundwater levels in immediate riparian zone.
One long and probably several short
peaks following main period of winter–
spring flooding.
Not known how long vigour is maintained
without flooding
River cooba
(Acacia
stenophylla)
1 in 3- 7 years
Not known. Seedlings possibly tolerant
of temporary waterlogging but duration
not known.
Not known, possibly maintains vigour for
up to 5 years without flooding. Trees near
creeks and waterbodies maintain vigour
much longer, possibly 10-15 years.
Small shrubs can
tolerate 1 in 7-10
years
2-3 months
Not likely to be
important
11
Species
Maintenance
Regeneration
Critical interval
Flood frequency
Flood duration
Timing of flooding
Coolibah
(Eucalytus
coolabah)
1 in 10-20 years;
drought hardy
Not known (water-logging is likely to
be detrimental)
Not expected to be
important. May be
important for
understorey plants.
Germination most likely on wet soils,
either following flood recession or in
run-on areas after rainfall.
Uncertain. Can maintain fair to good
condition for several years with no
flooding, being reliant on rainfall and
groundwater, possibly for 10-20 years
Cane Grass
(Eragrostis
australasica
1 in 2-3 years; will
tolerate 1 in 5-7
years
1-6 months
Non-critical
Nothing known about regeneration from
seed, seedling establishment or
circumstances when this is important.
Uncertain. Stems die off in less than a
year, but rootstock is assumed to persist
longer, possibly a few to several years.
Flooding to replenish seed bank is needed
at about 7 years.
Common reed
(Phragmites
australis)
1 in 1-2 years
8-12 months
Spring to autumn
Regeneration from rhizome most
important. Seeds commonly infertile or
low viability.
Reflood after 2-3 years to maintain vigour.
Can recover from up to 7 years without
flooding.
Water couch
(Paspalum
distichum)
1 in 1-2 years
5-8 months
Critical: late winter
or spring. Flooding
needed over
summer.
Regeneration from seed, not known. In
most instances, regeneration is
probably from rootstock.
Reflood after 2-3 years to maintain vigour.
Seeds short-lived, to 2 years, so seed
bank needs to be replenished almost
annually for regeneration from seed.
Rootstock persists 5-7 years in heavy clay.
Cumbungi
(Typha
domingensis and
T. orientalis)
Annual. Every 2-3
years may be
tolerable
8-12 months
Start in autumn–
winter. Dry phase
late summer into
autumn
Germination and early seedling growth
is on wet muds or shallow water.
Regeneration is any time from spring to
autumn.
Reflood after 2 years to maintain vigour,
but can recover from up to 5 years without
flooding
Marsh clubrush
(Bolboschoenus
fluviatilis)
Annual
3-5 months
Critical. Flooding to
start in late winter if
shoots are to
complete life cycle.
Regeneration from seed possibly not
important: may be reliant on regrowth
from rhizome and tubers.
Not certain. Reflood at about 3-5 years to
maintain vigour, but flooding needs to be
optimal to encourage recovery. May
recover after 5-7 years from rhizome and
tubers, but likely to be much less vigorous.
6 months is tolerable, if flooded
annually,
12
Table 4 Expected areas of inundation for selected flow volumes in the Macquarie Marshes
(based on Bowen and Simpson 2009 and NSW Department of Environment, Climate
Change and Water 2010d)
Flow volume (GL)
over 5 successive
months JuneApril/May at
Marebone weir
Area of floodplain
inundated (ha)
Area of common reed,
mixed marsh, water
couch and cumbungi
communities inundated
(ha)
Area of river
cooba and
lignum
communities
inundated (ha)
Area of river red
gum communities
inundated (ha)
100
19,000
7,744
477
9,705
250
50,000
13,395
1,728
23,437
400
80,500
16,325
2,353
29,674
700
145,160
19,884
2,890
35,526
Coolibah and black box woodlands are generally found in the Marshes on the less frequently flooded
parts of the floodplain. As a result, the NSW Department of Environment, Climate Change and Water
(2010c) included these with a range of flood tolerant communities in a functional group it called
‘floodplain vegetation’. For the four selected flow volumes the inundation extents for floodplain
vegetation varied between 1,400 ha and 75,000 ha.
Given that Bowen and Simpson (2009) mapped 8,412 ha of coolibah woodland and 16,114 ha of
black box woodland, MDBA has assumed that most of these communities will be inundated by the
700 GL flood volume. Analysis of modelled without-development flows between 1895 and 2009
show that the flow volumes selected from those determined by the NSW Department of
Environment, Climate Change and Water (2010c) would provide sufficient inundation frequency to
ensure the resilience of most flood-dependent vegetation in the Macquarie Marshes. For this
reason, these flows form the basis for the environmental water requirements for the Macquarie
Marshes.
Table 5 outlines the proposed flow indicators for vegetation communities of the Marshes. To
maintain semi-permanent wetlands and other lower elevation vegetation communities (including
some river red gum forest) a volume of 100 GL over a period of 5 months is proposed. To inundate a
larger proportion of the marshes, including the majority of river red gum forest and wetland
communities a volume of 250 GL over a period of 5 months is proposed. To inundate the broader
Marshes, including woodland communities, volumes of 400 GL and 700 GL over periods of 7 and 8
months respectively are proposed. The timing of these flows should be between June to April or
May to align with natural high flow periods.
5.2.2
Waterbirds
The Macquarie Marshes are renowned for supporting some of Australia’s largest waterbird breeding
events. The Macquarie Marshes Water Management Plan 1996 (NSW National Parks and Wildlife
Service & Department of Land and Water Conservation 1996), work undertaken by Kingsford and
Auld (2005), and the draft report on the ecological character of the Macquarie Marshes Nature
13
Reserve Ramsar site (NSW Department of Environment and Climate Change 2009b) link flood size
and duration to the size of breeding events for waterbirds.
The Macquarie Marshes Water Management Plan 1996 (NSW National Parks and Wildlife Service &
Department of Land and Water Conservation 1996) indicates that a flood of 250 GL may result in the
smallest number of breeding pairs of waterbirds at the fewest sites. For example, in 1993/94 flood
of 220 GL in 7 months enabled 4,600 pairs of intermediate egrets to successfully complete breeding.
At flows below this threshold, the area and duration of inundation might not be sufficient to support
a successful breeding event. As the volume of water increases above this threshold, there is a sharp
increase in the number of birds breeding. For instance, in 1990 when the water volume over a
seven-month period was 485 GL, there were 17,200 pairs of intermediate egrets and 65,000 pairs of
ibis breeding in the Marshes (NSW National Parks and Wildlife Service & Department of Land and
Water Conservation 1996). The Plan also noted that breeding starts no earlier than August, and has
not been recorded starting later than January.
Kingsford and Thomas (1995) found annual flows, measured at the Oxley gauge on the Macquarie
River, are significantly related to total colony size (number of nests) of waterbird species, including
intermediate egret, rufous night heron, glossy ibis, straw-necked ibis, Australian white ibis and royal
spoonbill. Analysis of breeding data between 1986 and 2001 indicates significant relationships
between numbers of colonies established and flow and flooded area. It also indicates that the best
predictor of nest numbers for all species is the amount of water flowing past Oxley in the three
months before breeding, although the strength of this relationship varies among species (Kingsford
and Thomas 1995; Kingsford and Johnson 1998; Kingsford and Auld 2005). Between 1978 and 2000,
colonial nesting waterbird breeding events commenced in the Marshes once inflow volumes
exceeded 200 GL (based on flow measured at the Oxley gauge), and the size of breeding events
increased with larger inflow volumes (Kingsford and Thomas 1995; Kingsford and Johnson 1998;
Kingsford and Auld 2005).
The draft report on the ecological character description of the Macquarie Marshes Nature Reserve
Ramsar site (NSW Department of Environment and Climate Change 2009b) states that the minimum
flow requirement for successful colonial nesting waterbird breeding throughout the entire Marshes
is flooding of sufficient volume and duration to inundate colony sites and feeding areas for at least
five consecutive months between August and March. According to the report, this requires between
180 GL and 300 GL, depending on preceding conditions.
The preceding information indicates that an inflow volume of around 250 GL to 300 GL (measured at
Marebone Weir) enables successful waterbird breeding. On this basis three of the flow indicators
proposed for vegetation outcomes are also likely to provide suitable conditions for colonial-nesting
bird breeding. The timing of proposed flow indicators for vegetation also aligns broadly with the
timing of bird breeding events.
5.2.3 Native fish
There is still debate in the scientific literature as to the relative role of flooding to fish community
dynamics, and an understanding of the nature of ‘fish ecology’-‘river flow’ interactions is by no
means clear (Humphries et al. 1999, Mallen-Cooper and Stuart 2003, Graham and Harris 2004; King
14
et al. 2009). For example, it has been suggested that some fish species, such as golden perch and
silver perch, require flow pulses or floods for spawning i.e. flood recruitment hypothesis (Humphries
et al. 1999). This is partly supported by King et al. (2009) which suggests that flow is one
environmental variable, although not always the key environmental variable, identified explaining
the occurrence and abundance of spawning of golden perch, silver perch and Murray cod at BarmahMillewa Forest. Other factors such water temperature and day length, or the interaction of a range
of environmental variables including flow, are suggested to also be important for native fish
recruitment (King et al. 2009).
Notwithstanding the ongoing debate regarding the link between hydrology and fish ecology,
available evidence suggests that provision of flows that connect the river channel to the floodplain
(e.g. Beesley et al. 2011), as well as in-channel flow variability, are important to sustaining key
ecological features such as native fish populations. Flow indicators described herein for flood
dependent vegetation communities and waterbirds are expected to provide outcomes to support
life-cycle and habitat requirements of native fish including provision of cues for spawning and
migration and access to food sources.
5.2.4 Other biota
There is little in the way of studies in the Macquarie examining flow-ecology relationships with
regard to other faunal groups. Nevertheless, the MDBA is confident that the specified environmental
water requirements for floodplain wetlands and waterbirds will have valuable beneficial effects on
the life-cycle and habitat requirements of amphibians, and water-dependent reptiles and
invertebrates. Key ecosystem functions associated with river and floodplain connectivity will also be
enhanced.
5.2.5 Proposed flow indicators
The site-specific flow indicators for the Macquarie Marshes are set out in Table 5. Generally, the
flow indicator component with the greatest level of uncertainty across the Basin is the definition of
the desirable frequency of flows, expressed as the proportion of years an event is required. This
uncertainty is due to a number of reasons. Firstly, it is likely that there are thresholds for many
plants and animals beyond which their survival or ability to reproduce is lost, but the precise details
of those thresholds are mostly unknown or where there is information (for instance river red gum
communities) our knowledge is evolving. Secondly, vegetation communities are located across the
floodplain and would have experienced significant variability in their inundation frequency under
pre-development conditions which subsequently makes specification of a single frequency metric
deceptively certain. For many species and ecological communities the relationship between water
provisions and environmental outcomes may not be threshold based, rather there could be a linear
relationship between flow and the extent of environmental outcomes or the condition of a
particular ecological species/community.
Recognising the degree of confidence in specifying a desirable frequency, ‘low–uncertainty’ and
‘high–uncertainty’ frequency of flow events have been specified (Table 5). For the low–uncertainty
frequency, there is a high likelihood that the environmental objectives and targets will be achieved.
The lower boundary of the desired range is referred to here as the high uncertainty frequency. This
15
is effectively the best estimate of the threshold, based on current scientific understanding, which, if
not met, may lead to the loss of health or resilience of ecological communities, or the inability of
species to reproduce frequently enough to sustain populations. The high–uncertainty frequencies
attempt to define critical ecological thresholds. The high–uncertainty frequency is considered to
indicate a level beyond which the ecological targets may not be achieved.
For the Macquarie Marshes the proposed inundation frequencies for wetlands and vegetation
communities have been informed by the requirements of the dominant vegetation communities.
Current understanding of these requirements is set out in Table 3, adapted from Roberts and
Marston (2011).
For waterbird breeding, in the absence of detailed studies, the MDBA has used its judgement to
specify desired inundation frequencies for waterbird breeding that are consistent with the life cycle
requirements of bird species and fall between the frequencies experienced in the withoutdevelopment and current-arrangements model runs.
Two key factors dictate that waterbirds do not need to breed every year on the same river system
(Scott 1997). Firstly, Australian waterbirds are highly mobile and their mobility over large spatial
scales is a defining characteristic (Scott 1997; Overton et al. 2009). Most of the 80 odd species of
(non-vagrant) Murray-Darling Basin waterbirds that use inland wetlands have broad Australia-wide
distributions and it is believed that individuals of most species are capable of dispersing at the scale
of the continent (Overton et al. 2009). As such, prior to river regulation at least some individuals of
the more mobile waterbird species have would have been able to seek suitable conditions for
successfully breeding somewhere within the Basin in most years (Scott 1997).
Secondly, it is not essential for waterbirds to breed every year to maintain sustainable populations
as they are generally long-lived (Scott 1997). Waterbirds become sexually mature at the age of one
to two years and have a life expectancy ranging generally from 3-4 years for ducks, up to 8 years for
larger birds such as ibis (Scott 1997).
These two key factors have informed the frequency of events for site-specific flow indicators
intended to support the habitat requirements of waterbirds, including provision of conditions
conducive to successful breeding of colonial nesting waterbirds. Specifically, it is desirable to provide
multiple opportunities for successful waterbird breeding within the range of their life expectancy.
The proposed flow indicators are consistent with this rationale.
It is recognised that periods between inundation events are an important consideration when trying
to determine ecosystem resilience or thresholds of irreversible change. When investigating the
environmental water requirements for the various sites, consideration was given to specifying a
maximum period between events or metrics related to maximum dry. However, the literature
regarding the tolerance of various floodplain ecosystems to dry periods is limited. In addition where
this information exists, recommended maximum dry intervals often conflicts with the maximum dry
experienced under modelled without development conditions.
Considering these issues, MDBA has not proposed a maximum dry period with the exception of a
small number of sites across the Basin, which does not include the Macquarie Marshes. Even so, the
16
importance of maximum dry periods and their role in maintaining ecosystem resilience is
recognised. Maximum dry periods between successful events is reported for hydrological modelling
associated with the Macquarie Marshes indicator site (see MDBA 2012) despite reducing the
maximum period between events not being the primary objective of the modelling process.
17
Table 5 Site-specific ecological targets and associated flow indicators for Macquarie Marshes
Site-Specific Flow Indicators
Event
Frequency-proportion of years
event required to achieve target
(%)
Site-Specific Ecological Targets
Flow volume
required (GL)
Provide a flow regime which ensures the current
extent of native vegetation of floodplain and
wetland communities is sustained in a healthy,
dynamic and resilient condition
Provide a flow regime which supports the habitat
requirements of waterbirds and is conducive to
successful breeding of colonial nesting waterbirds
Provide a flow regime which supports recruitment
opportunities for a range of native aquatic species
(e.g. fish, frogs, turtles and invertebrates)
Provide a flow regime which supports key
ecosystem functions, particularly those related to
connectivity between the river and the floodplain.
Note:
Without-development and baseline event
frequencies
Timinga
Low
uncertainty
(%)
High
uncertainty
(%)
Proportion of
years event
occurred under
modelled withoutdevelopment
conditions (%)
Proportion of
years event
occurred under
modelled
baseline
conditions (%)
100
Volume to be provided with
5 successive months
between June and April.
85
80
91
80
250
Volume to be provided with
5 successive months
between June and April.
50
40
66
35
400
Volume to be provided within
7 successive months
between June and April
40
30
49
27
700
Volume to be provided within
8 successive months
between June and May
17
17
19
17
Multiplication of the flow by the frequency (proportion of years event required) does not translate into the additional volume of water the site needs to be
environmentally sustainable. This is because part of the required flow is already provided under baseline conditions. Additional environmental water required is the
amount over and above the baseline flows.
18
6. Flow delivery constraints
Basin wide environmental objectives have been developed within the context of being deliverable in
a working river system that contains public and private storages and developed floodplains. To
understand and assess the implications of key constraints on the ability to achieve flow indicators at
the Macquarie Marshes, MDBA has drawn upon a combination of existing information (e.g. Water
Sharing Plans, flood warning levels) and practical knowledge of river operators supported by testing
using hydrological modelling.
The watering requirements (and thus objectives) of Section 5 are met through an appropriate water
delivery regime. Implementation of a delivery regime is potentially subject to a number of
constraints that may mean that environmental requirements are not met at all times. An example of
the constraints that apply to water delivery to the Macquarie Marshes is given below:

Prolonged flows of more than about 4,000 ML/d at Marebone Weir will cause flooding of
Gradgery Lane. Under current operating practices high priority is given to minimising the
period that a flow of 4,000 ML/d at Marebone Weir is exceeded.
Recognising that the delivery of environmental flows is highly dependent on existing system
constraints, the site-specific flow indicators for the hydrologic indicator sites across the Basin have
been classified into three broad types (Table 6). Despite the delivery of environmental flows being
highly dependent on existing system constraints, the site-specific flow indicators for Macquarie
Marshes are considered to be deliverable as mostly regulated flows under current operating
conditions.
Table 6 Site-specific flow indicators for the Macquarie Marshes and effect of system constraints
Site-specific ecological targets
Site-specific flow indicators
Provide a flow regime which ensures the current extent of
native vegetation of floodplain and wetland communities is
sustained in a healthy, dynamic and resilient condition
Achieve a total in-flow volume of 100 GL during
June to April for 80% of years
Provide a flow regime which supports the habitat requirements
of waterbirds and is conducive to successful breeding of
colonial nesting waterbirds
Provide a flow regime which supports recruitment opportunities
for a range of native aquatic species (e.g. fish, frogs, turtles
and invertebrates)
Provide a flow regime which supports key ecosystem
functions, particularly those related to connectivity between the
river and the floodplain
Achieve a total in-flow volume of 250 GL during
June to April for 40% of years
Achieve a total in-flow volume of 400 GL during
June to April for 30% of years
Achieve a total in-flow volume of 700 GL during
June to May for 17% of years
19
Key for Table 6
Achievable under current operating conditions
Flow indicators highlighted in blue are considered deliverable as mostly regulated flows under current
operating conditions.
Achievable under some conditions (constraints limit delivery at some times)
Flow indicators highlighted in yellow are considered achievable when delivered in combination with
tributary inflows and/or unregulated flow events. They may not be achievable in every year or in
some circumstances, and the duration of flows may be limited to the duration of tributary inflows.
Difficult to influence achievement under most conditions (constraints limit delivery at most
times)
Flow indicators highlighted in brown require large flows that cannot be regulated by dams and it is not
expected that these flows can currently be influenced by river operators due to the river operating
constraints outlined above.
7. Summary and conclusion
The Macquarie Marshes is a key environmental asset within the Basin and is an important site for
the determination of the environmental water requirements of the Basin. MDBA has undertaken a
detailed eco-hydrological assessment of Macquarie Marshes environmental water requirements.
Specified flow indicators are indicative of a long-term flow regime required to enable the
achievement of site-specific ecological targets at Macquarie Marshes and for the broader river valley
and reach. Along with other site-specific flow indicators developed across the Basin at other
hydrologic indicator sites, these environmental flow requirements were integrated within
hydrological models to inform the ESLT. This process, including consideration of a range of
constraints such as the one outlined in Section 6, is described in further detail within the companion
report on the modelling process ‘Hydrologic modelling to inform the proposed Basin Plan: Methods
and results’ (MDBA 2012).
20
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Kingsford, RT & Johnson, WJ 1998, ‘Impact of water diversions on colonially nesting waterbirds in
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23
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24
Appendix A
Data used in producing hydrologic indicator site maps
Data
Dataset name
Sourcea
Basin Plan regions
Draft Basin Plan Areas 25 May 2010
Murray–Darling Basin Authority (2010)
Dam walls/barrages
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia 2006
Gauges
100120 Master AWRC Gauges
Icon sites
Living Murray Indicative Icon Site Boundaries
Murray–Darling Basin Commission
(2007)
Irrigation areas
Combined Irrigation Areas of Australia Dataset
Bureau of Rural Sciences (2008)
Lakes
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia (2006)
Maximum wetland
Wetlands GIS of the Murray–Darling Basin Series 2.0
Murray–Darling Basin Commission
extents
(Kingsford)
(1993)
National parks/nature
Digital Cadastral Database
New South Wales Department of
reserves
Lands (2007)
National parks/nature
Collaborative Australian Protected Areas Database —
Department of the Environment,
reserves
CAPAD 2004
Water, Heritage and the Arts (2004)
Nationally important
Directory of Important Wetlands in Australia Spatial
Department of the Environment,
wetlands
Database
Water, Heritage and the Arts (2001)
Ocean and landmass
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia (2006)
Ramsar sites
Ramsar wetlands in Australia
Department of the Environment,
Water, Heritage and the Arts (2009)
Rivers
Surface Hydrology (AUSHYDRO version 1-6)
Geoscience Australia (2010)
Roads
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia (2006)
State border
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia (2006)
State forests
Digital Cadastral Database
New South Wales Department of
Lands (2007)
Towns
GEODATA TOPO 250K Series 3 Topographic Data
Geoscience Australia (2006)
Weirs
Murray–Darling Basin Weir Information System
Murray–Darling Basin Commission
(2001)
Weirs 2
a
River Murray Water Main Structures
Murray–Darling Basin Authority (2008)
Agency listed is custodian of relevant dataset; year reflects currency of the data layer.
25
Appendix B
Species relevant to criteria 1 and 4: Macquarie Marshes
Species
Recognised in
international
agreement(s)1
Environment
Protection
and
Biodiversity
Conservatio
n Act 1999
(Cwlth)
Fisheries
Management
Act 2004
(NSW)
Threatened
species
conservation
Act 1995
(NSW)
Amphians and reptiles
Sloane’s froglet (Crinia sloanei)5
V
Birds
Australasian bittern (Botaurus poiciloptilus)2
V
Australian bustard (Ardeotis australis)2
E
Barking owl (Ninox connivens)2
V
Bar-tailed godwit (Limosa lapponica)2

Black-breasted buzzard (Hamirostra
V
melanosternon)2
Black-chinned honeyeater (eastern subspecies)
V
(Melithreptus gularis gularis)2
Black-necked stork (Ephippiorhynchus asiaticus)2
E
Black-tailed godwit (Limosa limosa)2, 3
V
Blue-billed duck (Oxyura australis)2
V
Brolga (Grus rubicundus)
V
Brown treecreeper (Climacteris picumnus)2
V
Bush stone-curlew (Burhinus grallarius)2
E
Caspian tern (Hydroprogne caspia)2, 3

Cattle egret (Ardea ibis)2, 3

Common greenshank (Tringa nebularia)2

Common sandpiper (Actitis hyoleucos)2

Cotton pygmy goose (Nettapus coromandelianus)2
Curlew sandpiper (Calidris ferruginea)2
Diamond firetail (Stagonopleura guttata)2
E

V
26
Species
Eastern great egret (Ardea modesta)2, 3
Recognised in
international
agreement(s)1
Environment
Protection
and
Biodiversity
Conservatio
n Act 1999
(Cwlth)
Fisheries
Management
Act 2004
(NSW)
Threatened
species
conservation
Act 1995
(NSW)

Freckled duck (Stictonetta naevosa)2
V
Glossy black-cockatoo (Calyptorhynchus lathami)2
V
Glossy ibis (Plegadis falcinellus)2, 3

Grey-crowned babbler (Pomatostomus temporalis)2
V
Hooded robin (Melanodryas cucullata)2
V
Latham’s snipe (Gallinago hardwickii)2, 3

Magpie goose (Anseranas semipalmata)2
V
Major Mitchell’s cockatoo (pink cockatoo)
V
(Lophochroa leadbeateri)2
Marsh sandpiper (Tringa stagnatilis)2

Masked owl (Tyto novaehollandiae)5
V
Osprey (Pandion haliaetus)2
V
Painted honeyeater (Grantiella picta)2
V
Painted snipe (Rostratula benghalensis)
V
E
Red-backed button-quail (Turnix maculosa)2
V
V
Red-necked stint (Calidris ruficollis)2

Red-tailed black-cockatoo (Calyptorhynchus
V
banksii)2
Sharp-tailed sandpiper (Calidris acuminata)2, 3

Square-tailed kite (Lophoictinia isura)2
V
Superb parrot (Polytelis swainsonii)2
V
Turquoise parrot (Neophema pulchella)2
V
V
White-bellied sea-eagle (Haliaeetus luecogaster)3

Wood sandpiper (Tringa glareola)2

Fish
Murray cod (Maccullochella peelii peelii)2
V
27
Species
Recognised in
international
agreement(s)1
Environment
Protection
and
Biodiversity
Conservatio
n Act 1999
(Cwlth)
Silver perch (Bidyanus bidyanus)2
Fisheries
Management
Act 2004
(NSW)
Threatened
species
conservation
Act 1995
(NSW)
V
Mammals
Little pied bat (Chalinolobus picatus)2
V
Squirrel glider (Petaurus norfolcensis)2
V
Yellow-bellied sheathtail bat (Saccolaimus
V
flaviventris)2
Koala (Phascolarctos cinereus)5
V
Eastern freetail bat (Mormopterus norfolkensis)2
V
Stripe-faced dunnart (Sminthopsis macroura)2
V
Plants
Aromatic pepper-cress (Lepidium hyssopifolia)2
E
Rock fern (Cheilanthes sieberi subsp.
E
pseudovellea)5
Greenhood orchid (Pterostylis cobarensis)5
V
Pine donkey orchid (Diuris tricolor)5
V
Red Darling pea (Swainsona plagiotropis)5
V
Spiny mint-bush (Prostanthera spinosa)5
V
Communities
Aquatic ecological community of the Macquarie
E
Marshes4
Coolibah – black box woodland of the northern
Riverine Plains in the Darling Riverine Plains and
Brigalow Belt South bioregions
E
4
Myall Woodland in the Darling Riverine Plains,
Brigalow Belt South, Cobar Peneplain, Murray–
E
Darling Depression, Riverina and NSW South
Western Slopes bioregions4
28
E = endangered V = vulnerable
1 Japan–Australia Migratory Bird Agreement, China–Australia Migratory Bird Agreement, or Republic of
Korea – Australia Migratory Bird Agreement
2 NSW Department of Environment, Climate Change and Water (2009a)
3 NSW Department of Environment and Conservation (2006)
4 NSW Department of Environment, Climate Change and Water (2009b)
5 NSW Department of Environment, Climate Change and Water (2009a)
29